Method for removal of ammonia and related contaminants from water

ABSTRACT

A sono-molecular-conversion device and method for treating waste water including (a) feeding the waste water containing organic matter through a first sono-molecular conversion device including a plurality of ultrasound transducers; (b) applying ultrasonic energy to the waste water containing the organic matter by the sono-molecular conversion device to ultrasonically collapse microsized bubbles with transient cavitation in said waste water containing organic matter to effect mineralization of the organic matter into ammonia therein by sono-molecular-conversion; (c) feeding the waste water containing the ammonia through a second sono-molecular conversion device including a plurality of ultrasound transducers; and (d) applying ultrasonic energy to the waste water containing the ammonia by the sono-molecular conversion device to ultrasonically collapse microsized bubbles with transient cavitation in said waste water containing the ammonia to effect nitrification of the ammonia into nitrates and nitrites therein by sono-molecular-conversion.

CROSS-REFERENCE TO RELATED APPLICATIONS

The present application is a continuation in part of U.S. Ser. No. 12/588,543, filed on Oct. 19, 2009. U.S. Ser. No. 12/588,543 is a continuation-in-part of U.S. Ser. No. 11/534,008, filed on Sep. 21, 2006 now U.S. Pat. No. 7,624,703, which claims the benefit under 35 USC 119(e) of U.S. Provisional Patent Application No. 60/719,616, filed Sep. 22, 2005. U.S. Ser. No. 11/534,008 is a continuation-in-part of U.S. Ser. No. 11/042,607, filed in the U.S. on Jan. 25, 2005 now U.S. Pat No. 7,393,323. The subject matter of U.S. Provisional Patent Application No. 60/719,616; U.S. Ser. Nos. 12/588,543; 11/534,008; and 11/042,607 is incorporated herein by reference.

FIELD OF THE INVENTION

This invention relates to a non-microbial method and device for detoxification of ammonia, nitrite and nitrates by nitrification and mineralization of carbon suspended solids contained by water, including, but not limited to tertiary waste water intended for discharge into public waterways and lakes by petroleum processors, paper-makers, and steel manufacturers, among others. It also relates to treatment of phosphoric acid, lignin, and cellulose.

BACKGROUND OF THE INVENTION

McMaster University Centre for Engineering and Public Policy brought to public notice an Apr. 29, 2010, “Climate of Change” Symposium: “Making the Lakes Great”. The stated objectives are discussions on actions which will affect Ecosystem Threat Reduction and thereby adapt or improve resilience of the large lakes and also mitigate green house gas emissions and effect.

The present application includes process separation between the nitrification, and mineralization for providing continuous, environment-friendly nitrogen (N₂) release. Although nitrogen (N₂) release is possible with current microbial de-nitrification, it could prove unsatisfactory for addressing the vast quantity of global industrial waste water at hand and curbing global warming because of its necessary release of carbon dioxide and methane green house gases to atmosphere.

U.S. Ser. No. 11/534,008 discloses non-microbial ammonia reduction with continuous recirculation contaminant flow where an accumulating rate (mg/l/hr) of fish generated ammonia concentration was negated by an opposite and opposing rate of sonic ammonia molecular dissociation.

Contaminated tertiary waste water, delivered by industry for de-contamination contains significant ammonia or nitrate concentrations which can be reduced to an acceptable regulatory level with either a SMC (sono-molecular conversion) low-volume single molecular dissociation pass, or a high volume with repetitive recirculation molecular dissociation passes.

At a specific rate (mg/l/hr), this disclosure relates to associating nitrate/nitrite to ammonia while mineralizing organic carbon to ammonia (NH₃), thereafter, nitrification, dissociates NH₃ to nitrite (NO₂), then dissociates nitrite to nitrate (NO₃) and finally dissociates nitrate to nitrogen gas (N₂) where after the de-contaminated tertiary waste water is ready for discharge into public waterways and/or Great Lakes.

Current microbial processing technology for treating industrial tertiary waste water ammonia consists of two separate microbial processes; the first for ammonia nitrification and the second for nitrate de-nitrification. The device name applied to these two waste water treatment processes is “Sequencing Batch Reactor” (SBR).

For the nitrification-only purposes, the reactor is tagged single-stage and for de-nitrification-only purpose, second-stage.

The Single Stage Reactor performs an aerobic bacteria nitrification process, changing ammonia (NH₃) to nitrite (NO₂), and then the nitrite to nitrate (NO₃). After that, the nitrate (NO₃) is transferred into the Second Stage Reactor along with added organic carbon, such as methanol, thereby providing an anoxic substrate for aerobic/anaerobic bacteria to denitrify nitrate (NO₃) into nitrogen (N₂) gas for atmospheric release. Unfortunately, in performing the conversions, these same bacteria generate carbon dioxide (CO₂) and methane (CH₄), which is released into the atmosphere as green house gas.

The role of nitrosomonas, nitrobacter and heterotrophic bacteria resident in a bio filter is highlighted by Steven T. Summerfelt and Mark J. Sharrer of CFFI, who discuss nitrification and de-nitrification bacteria generating CO₂.

When ammonia is added to water a large percentage combines with the water molecules forming a combined substance called Ammonium. Ammonia combined this way with water is called NH₄ N and is ionized, while that which does not combine with water is called non-ionized NH₃ N. The ratio between the two substances varies with water pH. When pH is high, say 9, the percentage of NH₃ is high vs. NH₄, and if pH is 6, NH₄ is high vs. NH₃. A large fraction of CO₂ is produced by the nitrification bacteria in the bio filter as they consume 4.6 mg/l of oxygen while producing 5.9 mg/l of CO₂ for every 1 mg/l of TAN (NH₃ N+NH₄ N) consumed and the heterotrophic bacteria another 1.38 mg/l of CO₂ for every 1 mg/l of DO used by nitrification bacteria.

OBJECTS AND SUMMARY

An object of this invention is to provide an improved method and apparatus for eliminating ammonia and reducing nitrite and nitrate and organic carbon concentrations present in industrial tertiary waste-water.

An object of this invention is replacement of bacterial oxidation by the science of matter, the branch of natural sciences dealing with the composition of substances, their properties, associations and dissociations. Dissociation, usually reversible, (association), is a field of science where action of high temperature and pressure causes molecules to split into simpler groups of atoms, single atoms or ions.

According to one embodiment, a sono-molecular-conversion method for effecting nitrification of ammonia in water comprises feeding the water containing ammonia through a sono-molecular conversion device including a plurality of ultrasound transducers, and applying ultrasonic energy to the water containing ammonia by the sono-molecular conversion device to ultrasonically collapse microsized bubbles with transient cavitation in said water containing ammonia to effect nitrification of ammonia therein by sono-molecular-conversion.

This disclosure is based on the considerable research by the inventor in the field of low-frequency ultrasound with respect to implosive transient cavitations bubble collapse wherein the very high temperatures (5,000° K.) and pressures (500 atmospheres) caused nitrification through dissociation of ammonia (NH₃) to nitrite (NO₂) and nitrite (NO₂) to nitrate (NO₃) and nitrate (NO₃) to nitrogen gas (N₂+2H₂O+1/2O₂).

Another embodiment of this invention relates to mineralization wherein very high temperatures and pressures in conjunction with organic carbon (CH₃) or (CH₄) caused association where nitrate (NO₃) was reverted to nitrite (NO₂) and nitrite (NO₂) was reverted to ammonia (NH₃).

Another embodiment of this disclosure is that mineralization and nitrification is made possible at any frequency of ultrasound that transient cavitations bubble collapse induces the necessary high temperature and pressure.

Another embodiment of this disclosure relates to suspended-solids ultrasonic pulverization which provides a suspended, uninterruptible micron sized inorganic particle flow.

Another embodiment of this disclosure relates to release of aqueous entrained anoxic gas (N₂) for atmospheric dispersal.

BRIEF DESCRIPTIONS OF DRAWINGS

FIGS. 1A through 1D illustrates views of a self-contained, SMC console containing the components necessary to decontaminate industrial tertiary waste water in-flow according to an embodiment of the present invention.

FIG. 2 illustrates a sono-molecular conversion device according to one or more embodiments of the present invention.

FIG. 3 is a chart showing ammonia nitrification at 2 W/cm².

FIG. 4 is a chart showing ammonia nitrification at 1 W/cm².

FIG. 5 is another chart showing ammonia nitrification.

FIG. 6 is a chart showing ammonia mineralization at 80 W/cm².

FIG. 7 is another chart showing ammonia nitrification at 80 W/cm².

FIG. 8 is a schematic diagram of an embodiment of the invention useful for waste water treatment.

FIG. 9 is a diagram of a conventional pipe system.

DETAILED DESCRIPTION OF THE PREFERRED EMBODIMENTS

A major technological difference between a bio filter and the sono molecular-conversion processes is that the former relies upon bacterial digestive oxidation processes of living aerobic and anaerobic organisms while the latter relies upon the science of matter, where high temperature and pressure initiates molecular dissociation and association causing molecules to split into simpler groups of atoms, single atoms or ions.

Sono-Molecular-Conversion Nitrification (Dissociation):

The inventor's experimentation, has demonstrated the following interrelationships associated with sono-molecular-conversion nitrification (dissociation) of ammonia (NH₄/NH₃). Ammonia/water mixtures were irradiated with ultrasound pressure waves having a frequency of 30 kHz and intensity settings of 2.0, 1.5, and 1.0 W/cm². The corresponding pressure amplitudes were, respectively, 212 kPa, 150 kPa, and 100 kPa. The ammonia/water concentrations were 2.0, 4.0, 8.0, and 250 mg/L. The water sources, variably experimented with, were municipal, spring and distilled.

FIGS. 3 and 4 and the following tables illustrate the results of the experiments:

EXPERIMENT # 1 - Nitrification (Dissociation) Results Summary Table - (see FIG. 3) Status pH DO NH₄/NH₃ NO₂ NO³ INTENSITY TIME Start 7.6 9.5 mg/l 2 mg/l   0 mg/l <5 mg/l 2 W/cm²  0 Hrs Finish 7.6 9.5 mg/l 0 mg/l <0.5 mg/l 10 mg/l 2 W/cm² 21 Hrs

EXPERIMENT # 2 - Nitrification (Dissociation) Result Summary Table - (see FIG. 3) Status pH DO NH₄/NH₃ NO₂ NO₃ INTENSITY TIME Start 7.6 10 mg/l 4 mg/l    0 mg/l  5 mg/l 2 W/cm²   0 Hrs Finish 7.6  8 mg/l 0 mg/l <0.25 mg/l 10 mg/l 2 W/cm² 20.5 Hrs

EXPERIMENT # 3 - Nitrification (Dissociation) Results Summary Table - (see FIG. 3) Status pH DO NH₄/NH₃ NO₂ NO₃ INTENSITY TIME Start 7.6 9.5 mg/l 8 mg/l    0 mg/l  5 mg/l 2 W/cm²   0 Hrs Finish 7.6 9.5 mg/l 0 mg/l <0.25 mg/l 10 mg/l 2 W/cm² 20.5 Hrs

EXPERIMENT # 4 - Nitrification (Dissociation) Results Summary Table - (see FIG. 3) Status pH DO NH₄/NH₃ NO₂ NO₃ INTENSITY TIME Start 7.6 9.5 mg/l 250 mg/l    0 mg/l  5 mg/l 2 W/cm²  0 Hrs Finish 7.6 9.0 mg/l  0 mg/l <0.25 mgl >5 mg/l 2 W/cm² 20 Hrs

EXPERIMENT # 5 - Nitrification (Dissociation) Results Summary Table - (see FIG. 4) Status pH DO NH₄/NH₃ NO₂ NO₃ INTENSITY TIME Start 7.6 9.5 mg/l 4 mg/l   0 mg/l  5 mg/l 1 W/cm²  0 Hrs Finish 7.6  10 mg/l 0 mg/l 0.25 mg/l 10 mg/l 1 W/cm² 40 Hrs

The following observations were made as a result of the experiments:

1) For equal water volumes containing different concentrations of ammonia, the time required to reduce all such varying ammonia concentrations to zero was the same.

2) The time required to decrease a given total ammonia concentration in water to zero was inversely proportional to the applied sono-molecular-conversion intensity, (W/cm²). For example, the time necessary to bring total ammonia concentration in water to zero with an applied sono-molecular-conversion intensity of 2 W/cm² was half that required at 1 W/cm².

3) After sono-molecular-conversion irradiation reduced total ammonia concentration in water to zero, the remaining residual concentrations of nitrite and nitrate remained unchanged with continuing sono-molecular-conversion irradiation. Further, at this point, even with several sequentially added ammonia concentrations being reduced to zero by sono-molecular-conversion, the residual concentrations of nitrite and nitrate showed only slight increase.

4) Following initial nitrification, the residual concentration of nitrite was 0.25 mg/L and the residual concentration of nitrate was 5 mg/L.

5) Following each sono-molecular-conversion, nitrification (dissociation) experiment, water pH remained virtually unchanged, i.e., the increase in pH was slight. After each sono-molecular-conversion experiment was completed, the concentration of dissolved oxygen remained the same or showed a slight increase.

6) The above sono-molecular-conversion nitrification (dissociation) experiment results were independent of temperature of the water/ammonia mixture over the range of 48° F. to 87° F.

For the above experiments, an 8.5 liter experimental tank volume contained 8,421,000 mg of water. The ammonia concentrations employed were 2 mg/l, 4 mg/l, 8 mg/l and 250 mg/l. Therefore, the corresponding weight of ammonia was 17 mg, 34 mg, 68 mg and 2125 mg, and the % weight of ammonia in tank water was 0.0002%, 0.0004% 0.0008% and 0.025%.

Water and ammonia molecules weigh the same on the chemical scale. A water molecule consists of 2 atoms of hydrogen and 1 atom of oxygen while an ammonia molecule consists of 1 atom of nitrogen and 3 atoms of hydrogen. When ammonia is added to water having a pH of 7, 99% of the ammonia molecules bond with water molecules forming ammonium (NH₄) ions. Ammonium ions repel one another. Ammonia (NH₃) is polar and as such readily dissolves in water.

The end result is establishment of a widely separated 3D lattice-work of ammonium ions submerged within the experimental tank water volume. Within the experimental tank water is a seemingly endless invisible fog of micron size contaminant nucleation sites interspersed relatively evenly throughout the water volume. When ultrasonic irradiation commences, a significant number of nucleation sites will form micron size bubbles which, with each succeeding pressure wave, will grow until they finally collapse. This cavitations process is repeated over and over again while ultrasonic irradiation continues. However, since the population of ammonium ions is evenly distributed throughout the water volume, there is an equal chance that the ammonium ion population particular to each ammonia/water concentration will experience the same percentage loss of ammonium ions to nitrification at the same time.

Hence, all the above levels of ammonia/water concentrations will, as the experiment confirmed, complete the reduction of ammonia concentration to zero in the same time period as each curve is asymptotic to zero.

It was reported by O. I. Babikov in 1960, that increasing ultrasonic intensity (W/cm²) shortened the time from cavitations bubble initiation to its catastrophic collapse. More precisely, it is an increase in both the rare factional and compressive pressure wave amplitudes that shortens the time from cavitations bubble initiation to its catastrophic collapse. Therefore, increasing the ultrasonic pressure amplitude increases the frequency of all individual micro sized bubble initiation to collapse events than will occur at lower ultrasonic pressure amplitudes. Since each ammonium ion situated adjacent to a collapsing micro sized bubble undergoes the nitrification process it follows that increasing ultrasonic pressure amplitude shortens the time to reduce a given ammonia/water concentration to zero. FIG. 7 demonstrates the relationship between ultrasonic pressure amplitude and the sono-molecular-conversion-process duration, in hours, necessary to reduce all the above ammonia/water concentrations to zero.

Sono-Molecular-Conversion Mineralization:

The inventor also experimented with sono-molecular-conversion of organic waste (uneaten fish-food) into inorganic ammonia. The fish-food/water mixtures were irradiated at an ultrasound frequency of 30 kHz at intensity settings of 2.0 and 1.0 W/cm². The concentration of fish food was 1.1 gm/L. The water source experimented with was municipal.

FIGS. 3 and 4 and the following tables illustrate the results of the experiments.

EXPERIMENT # 6 - Mineralization Results Summary Table (TETRAFIN flakes, 0.38 gm/l), (see FIG. 6) Denitrification (Association) pH DO NH₄/NH₃ NO₂ NO₃ INTENSITY TIME Start 7.4 9.5 mg/l 0 mg/l 0.25 mg/l   5 mg/l 2 W/cm² 0 Hrs Finish 0.5 mg/l   0 mg/l 0 mg/l 2 W/cm² 3 Hrs Mineralization Start 0.5 mg/l   0 mg/l 0 mg/l 2 W/cm² 3 Hrs Finish 4 mg/l 0 mg/l 0 mg/l 2 W/cm² 7 Hrs Nitrification (Dissociation) Start 4 mg/l 0 mg/l 0 mg/l 2 W/cm² 7 Hrs Finish 7.4 9.5 mg/l 0 mg/l 0.25 mg/l   5 mg/l 2 W/cm² 35 Hrs 

EXPERIMENT #7 - Mineralization Results Summary Table (CHICLID pellets, 0.38 gm/l), (see FIG. 6) Denitrification (Association) pH DO NH₄/NH₃ NO₂ NO₃ INTENSITY TIME Start 7.4 9.5 mg/l 0 mg/l 0.25 mg/l   5 mg/l 2 W/cm² 0 Hrs Finish 1 mg/l 0 mg/l 0 mg/l 2 W/cm² 2 Hrs Mineralization Start 1 mg/l 0 mg/l 0 mg/l 2 W/cm² 2 Hrs Finish 8 mg/l 0 mg/l 0 mg/l 2 W/cm² 9 Hrs Nitrification (Dissociation) Start 8 mg/l 0 mg/l 0 mg/l 2 W/cm² 9 Hrs Finish 7.4 9.5 mg/l 0 mg/l <0.25 mg/l    5 mg/l 2 W/cm² 42 Hrs 

The inventor's experimentation demonstrated the following interrelationships applicable to sono-molecular-conversion of organic fish waste (uneaten fish-food) into inorganic ammonia.

1) For equal water volumes containing the same measure of organic matter, (fish-food), the time required to reduce organic matter to zero was the same. Zero Organic Matter Concentration was defined as the level of highest ammonia concentration converted by the mineralization process.

2) The time required to decrease a given organic matter concentration to zero (as defined in 1, above) was inversely proportional to the applied ultrasonic intensity (W/cm²). For example, the time necessary to bring organic matter concentration in water to zero with an applied ultrasonic intensity of 2.0 W/cm² was half that required at 1.0 W/cm².

3) Following each sono-molecular-conversion mineralization experiment, the water pH remained virtually unchanged, i.e., the increase in pH was slight. After each sono-molecular-conversion mineralization experiment was completed the concentration of dissolved oxygen remained the same or showed a slight increase.

4) Coincident with the point of peak ammonia concentration and the simultaneous reduction of carbon to zero, the nitrification process automatically resumed and continued until the ammonia was reduced to 0.0 mg/L.

Sono-Molecular-Conversion Denitrification (Association):

The inventor's experimentation, demonstrated the following interrelationships are applicable to sono-molecular-conversion denitrification (association) and occurred concurrently with the mineralization conversion of organic matter (uneaten fish-food) to inorganic ammonia.

1) Before denitrification (association), the residual concentration of nitrite in water was <0.25 mg/L and the residual concentration of nitrate was 5 mg/L.

2) Very rapidly following the sono-molecular-conversion initiation of the mineralization process, the above nitrite and nitrate concentrations within the aqueous medium were converted to NH₃.

3) Thereafter, nitrite and nitrate concentration remained at 0.0 mg/L throughout the mineralization process, i.e., until the concentration of carbon was exhausted and ammonia concentration had peaked.

4) For equal water volumes containing the same measure of organic matter (uneaten fish-food), the time required to decrease a given residual concentration of nitrite and nitrate to zero was the same.

5) The time to decrease a given concentration of nitrite and nitrate to zero was inversely proportional to applied sono-molecular-conversion intensity (W/cm²).

For example, the time necessary to bring nitrite and nitrate concentration in water to zero with a sono-molecular-conversion intensity of 2.0 W/cm² was half the time required at 1.0 W/cm².

6) Following each sono-molecular-conversion nitrification (association) experiment, the water pH remained virtually unchanged, i.e., the increase in pH was slight. After each sono-molecular-conversion nitrification (association) experiment was completed, the concentration of dissolved oxygen remained unchanged or showed a slight increase.

Sono-Molecular-Conversion Nitrification/Mineralization/Denitrification:

Each of the above water/contaminate mixture experiments were conducted separately using discrete but varying measures of ammonia (NH₃) and organic fish food.

Nitrification (Dissociation):

Several separate concentrations of NH₃ were added to the same, but separate volumes of water. Such mixtures were irradiated at specific sono-molecular-conversion intensities (W/cm²) and with 30 kHz ultrasound to create continuous transient cavitations within the mixture until the NH₄/NH₃ concentration was reduced to 0.0 mg/L.

Mineralization:

Similarly, several concentrations of organic fish-food were added to the same, but separate volumes of water. Such mixtures were irradiated at specific sono-molecular-conversion intensities (W/cm²) and with 30 kHz ultrasound to create continuous transient cavitations within the mixtures until the organic (carbon) matter was fully converted into inorganic matter as indicated by the maximum concentration of ammonia converted.

Denitrification (Association):

Concurrent with the reduction of organic matter into inorganic matter (mineralization) it was observed that residual concentrations of nitrite (NO₂) and nitrate (NO₃) existing in the water volumes before commencement of the mineralization experiment were rapidly reduced to 0.0 mg/L and remained so throughout the mineralization conversion of organic matter to inorganic matter.

The above separate experiment objectives are combinable and function together as one continuous 24/7 synergistic sono-molecular-conversion process to secure the above nitrification, mineralization and association objectives.

In practice, the sono-molecular-conversion intensity (W/cm²), is variably adjusted to the rate of ammonia concentration generated in a given aquaculture tank volume by the quantity of fish contained therein and the quantity of fish-food employed. That is, the sono-molecular-conversion intensity is adjusted in amplitude to reduce ammonia concentration at a rate equal to, or greater than, the combined rate at which the fish gill/urine, fish-food and fish feces are generating ammonia.

The prime-mover for sono-molecular-conversion (SMC), in the aqueous medium is the presence of negative and positive alternating pressure waves which create micro-sized vapor-bubbles which, commensurate with the applied sono-molecular-conversion frequency, collapse upon reaching resonant size by a phenomenon known as transient cavitations. In the fish aquaculture SMC application, frequencies of interest extend over the ultrasonic range 20 to 60 kHz with 30 kHz being the frequency of choice.

The range for the sono-molecular-conversion intensity setting is adjustable from zero to 10 W/cm², (zero to 387 kPa) which corresponds to safe ammonia concentration reduction rate for fish cultured at a density of 5 lb/ft³ and estimated uneaten feed of 1 gm/L.

The preferred ammonia detoxification apparatus for a Recirculating Aquaculture System (RAS) illustrated by U.S. patent application Ser. Nos. 10/676,061, 10/912,608 and 11/042,607 is incorporated herein by reference, and can be used herein. However, the invention's SMC technology is applicable as a “stand alone” ammonia detoxification device for an existing RAS, as well as for integration with municipal and industrial organic waste reduction/conversion applications. The technology is also applicable to removing ammonia from waste waters, such as tertiary industrial waste water.

FIGS. 1A-D are side, rear, plan, and front elevations, respectively, of a sono-molecular conversion apparatus 52 used in one or more embodiments of the present invention that are applicable to removing ammonia from waste waters, such as tertiary industrial waste water.

Incoming water, such as waste water containing ammonia, is input through input 22 with the assistance of a peristaltic pump 5. The incoming water flows up through a pipe 26 into a first sono-molecular converter (SMC) 1, a more detailed view of which can be seen in FIG. 2. After exiting from the top of SMC 1, the fluid passes through a horizontal pipe 28 into a second SMC 1′. The water exiting the second SMC 1′ travels through a pipe 25 and out through output 24.

As best seen in FIG. 1C, each SMC includes a plurality of transducers 20 arranged in a circular pattern about a top portion of the SMC. The number of transducers used will depend on the characteristics of the transducers and the intended applications. One of ordinary skill in the art will be able to determine the appropriate number. In one embodiment, eight transducers are used. In another embodiment, twenty-five transducers are used. In some embodiments, as many as fifty transducers can be used.

An ultrasonic generator 2 generates ultrasonic energy and supplies the energy to the transducers 20. A console 3 includes electronics for controlling the water quality probes 6, 7, 8, 9, 10, 11 and water quality indicators 12, 13, 14, 15, 16, and 17, illustrated in FIGS. 1B and 1D. A power supply 4 provides power to the various components of the sono-molecular conversion apparatus.

The sono-molecular converter 1 is illustrated in cross-section in FIG. 2. At the bottom of the SMC 1 is a first conduit 74 which functions as an inlet for the SMC 1. At a region 76, above the first conduit 74, the diameter, and thus volume, of the SMC 1 is increased. The plurality of transducers 20 are equally spaced in a semicircular manner at the top of the SMC 1. The transducers 20 are angled so as to input ultrasound energy in an overlapping manner, as illustrated in FIG. 2.

At the top center of the SMC 1 is a second conduit 72 that functions as an outlet for the SMC 1. Conduit 74 is a high velocity, low pressure inlet. Due to the divergent shape at region 76, upon reaching the transmitting faces of transducers 20 the waste water flow is at very low velocity and high pressure. Conduit 72 venturi shaped exit is the means for the waste water resuming high velocity and low pressure exit flow characteristics.”

In view of the fact that the SMC 1 has a larger diameter at the expanded region 76, water flowing through conduits 72, 74 is slowed down while it is resident in the center section 76, thus increasing the dwell time of the liquid within the SMC 1.

The SMC 1 comprises two sections; an upper section comprising a circular stainless steel machined casting and a coned shaped stainless steel lower section. The machined casting and cone shaped section are bolted together and water sealed with an “O” ring gasket to form 72, 74 and 76.

Each of the transducers 20 comprise four elements, 1) an upper section containing a non-reflective component, 2) a piezo crystal bonded to the non-reflective upper section, 3) a polished stainless steel body with a threaded hole through its center and whose body is epoxy-bonded to a polished surface on the stainless steel casting and 4) a threaded bolt which passes through 1) and 2) and through thread tightening 3, anchors 1), 2) and 3) to the assembly comprising 72, 74 and 76.

Also of importance is the location and arrangement of the ultrasonic transducers. Current sono chemical practice relies upon positioning ultrasonic transducers around the external periphery of existing piping. Often such transducers will be placed facing each other on opposite sides of a pipe, i.e., in juxtaposition, resulting in standing ultrasonic waves or wave cancellation with unreliable and unpredictable results. Such a state-of-the-art flow through technique is illustrated in FIG. 9, wherein a pipe 202 has a plurality of transducers 204 arranged facing each other on opposite sides of the pipe 202.

The placing of the ultrasonic transducers 20 in the same plane, equi-spaced in a circular pattern, at an inclined angled, as illustrated in FIGS. 1C and 2, and all operating at the same frequency from one ultrasonic power source, makes for focused ultrasonic intensity magnification without incurring pressure wave interference. The result therefore is predictable sono-molecular dissociation.

With regard to the embodiments illustrated in FIGS. 1 and 8, the exact processes occurring in the SMC depend on which input effluent constituents are mixed with the waste water.

When the input constituents are organic materials such as organic carbon (CH₃) or (CH₄) and nitrates (NO₃), the process associates the NO₃ to NH₃ and mineralizes the organic carbon into ammonia (NH₃). In this situation, mineralization is the dominant process. Whenever organic carbon exists, the SMC will first mineralize the organic material, i.e., dissociating it into inorganic ammonia. Once the organic carbon is exhausted the SMC will automatically revert to the practice of nitrification (dissociation) with the end result being N₂.

When the input constituent is nitrate (NO₃) only, the process nitrifies (dissociates) the nitrates (NO₃) to N₂.

When the input constituent is ammonia only, the ammonia is converted by nitrification (dissociation) into NO₃, then to N₂.

After the nitrification (dissociation) has been completed, the effluent may be routed to a jet-pump venturi to bring entrained N₂ gas out of solution for release to atmosphere. The effluent is then discharged in aqueous form for detoxified release as required.

FIG. 6 demonstrates that, at the point of organic carbon exhaustion, the transition from mineralization to nitrification (dissociation) is automatic.

FIG. 7 demonstrates that regardless of ammonia concentration, sono-molecular conversion nitrification (dissociation) will take place in the same time period. Unlike bacteria driven processes, sono-molecular conversion requires no oxygen, or alkali or acid addition for pH adjustment.

FIG. 8 shows a waste water plant 300 utilizing SMC. Influent from households and businesses is delivered through pipe 302. The influent is screened at bar screens 304, and the removed screenings are taken to a landfill. The screened influent is stored in the wet well 306, and pumped through a pump house 308 into pipe 310.

At a primary settling tank 312, skimmings and grease are removed and sent to the landfill. After settling, primary sludge is delivered to a cyclone degritter 314 in order to remove grit that is also sent to the landfill. After passing through the degritter 314, the remainder is delivered to a first SMC 316, where the organic material in the remainder is converted to ammonia. In addition, phosphoric acid in the remainder will be converted into phosphate ions (PO₄). It is also possible that some of the ammonia will be nitrified in the first SMC 316.

The ammonia is then conveyed through conduit 318 to a second SMC 320, where the ammonia, as well as suspended solids from the settling tank 312, are delivered. In the second SMC 320, nitrification of the ammonia is caused by dissociating the molecules into nitrites (NO₂) and nitrates (NO₃). The nitrites and nitrates are then converted to nitrogen gas (N₂) in water, which is delivered to disposal or recycling 330. In addition, any remaining organic matter in the water may be converted into ammonia, and any phosphoric acid in the remainder may be converted into phosphate ions (PO₄).

The water quality probes 6, 7, 8, 9, 10, 11 can be used to monitor the pH and ammonia content of the water in order to control the residence time in the SMCs and/or the ultrasound intensity.

Concurrent Processing of Phosphoric Acid and Ammonia:

Phosphoric acid (H₃PO₄) is used in fertilizer formulation, detergents and food flavoring. Phosphoric acid (H₂PO₄) is used as a plating to resist steel corrosion and as a component of lithium batteries. Phosphate or Orthophosphate anions (PO₄) have many scientific investigatory uses and its crystals have been used in optical applications. Orthophosphoric acid (H₃PO₄) is a polar molecule and therefore highly soluble in water. Triprotic means that the orthophosphoric acid molecule can dissociate up to three times (Wikipedia).

-   1) H₃PO₄+H₂O>H₃O+H₂PO₄ required dissociation constant pKa1=2.12 (pH) -   2) H₂PO₄+H₂O>H₃O+HPO₄ required dissociation constant pKa2=7.21 (pH) -   3) HPO₄+H₂O>H₃O+PO₄ required dissociation constant pKa3=12.67 (pH) -   After the first dissociation, H₂PO₄, the dihydrogen phosphate anion     is dominant. -   After the second dissociation, HPO₄, the hydrogen phosphate anion is     dominant. -   After the third dissociation, PO₄, the phosphate or orthophosphate     anion is dominant. -   Collectively these three anions are called orthophosphates.     For a total given acid solution, -   [A]=[H₃PO₄]+[H₂PO₄]+[HPO₄]+[PO₄] is the total number of milligrams     of pure H₃PO₄ which have been used to prepare one liter of the     aqueous solution.     The following table from Wikipedia shows the various     interrelationships:

[A] [H₃PO₄] [H₂PO₄] [HPO₄] [PO₄] mg/l pH % [A] % [A] % [A] % [A] 30960 1.08 91.7 8.29 6.2 × 10/−6  1.6 × 10/−17 3096 1.62 76.1 23.9 6.2 × 10/−5 5.55 × 10/−16 309.6 2.25 43.1 56.9 6.2 × 10/−4 2.33 × 10/−14 < .1^(st). Dissociation. 31 3.05 10.6 89.3 6.20 × 10/−3  1.48 × 10/−12 3.1 4.01 1.30 98.6 6.19 × 10/−2  1.34 × 10/−10 0.31 5.00 0.133 99.3 0.612 1.30 × 10/−8 0.031 5.97 1.34 × 10/−2 94.5 5.50 1.11 × 10/−6 0.0031 6.74 1.80 × 10/−3 74.5 25.5 3.02 × 10/−5 0.00003 7.00 8.24 × 10/−4 61.7 38.3 8.18 × 10/−5 > 2^(nd) Dissociation. Current Phosphoric Acid Concentration Reduction Practice for Waste Water:

The substrate used to remove orthophosphate is air-activated sludge which, after processing, is converted into dry-cakes and made available for use as fertilizer.

1) Biological—aerobic bacteria present in the air-activated sludge consume more orthophosphate than is needed for their existence and along with the consumed orthophosphate they are discarded along with the used sludge substrate. This biological oxidation process is not sufficiently efficient and therefore is used in conjunction with chemical precipitation of the aqueous sludge to increase overall orthophosphate removal efficiency.

2) Chemical Precipitation—Lime or iron derivatives are added progressively to adjust the pH of the aqueous sludge. If, for example, as shown in the above table, at the beginning of the precipitation process the phosphoric acid concentration shown was 30,960 mg/l at pH 1.08 then by adding lime to bring the aqueous sludge typically to a pH of 5 the original concentration will have been lowered to 0.31 mg/l with the corresponding percentage composition of H₃PO₄, H₂PO₄, HPO₄ and PO₄ as shown alongside by the above Table.

SMC Phosphoric Acid Concentration Reduction Practice for Waste Water:

SMC technology, as demonstrated by the experimental data herein for ammonia nitrification and organic mineralization, does not employ molecular oxidation or chemical precipitation. Instead, induced high temperature and pressure in the range of 5,000° K. and 500 atmospheres initiates flameless combustion to dissociate (modify) original molecule atomic structure to its simplest molecular form.

It follows that whatever the initial aqueous orthophosphate form; SMC will dissociate that structure to its simplest molecular structure, namely PO₄. From the above Table, PO₄ orthophosphate concentration in waste water is virtually non-existent. For municipal waste water (sewage) treatment the concentration of orthophosphate in raw sewage is in the range 4-16 mg/l. In a Point Source, such as a fertilizer manufacturing plant, the orthophosphate concentration in raw waste water is in the range 160-200 mg/l. The proposed 2012 EPA Regulation for orthophosphate concentration in waste water effluent discharge must be in the range 0.01-0.03 mg/l, or less.

SMC Lignin, Cellulose and Glucose Dissociation:

In the search for alternate fuels from domestic sources the demand for ethanol has steadily increased. The two basic sources are starch feed stocks or cellulose feed stocks. Cellulose materials typically are paper, cardboard, wood and fibrous plant material.

SMC will feature cellulose material which is less productive than starch based materials such as corn. In contrast to starch feed stocks, cellulose bio mass is less expensive and more abundant. However, it is the structural complexity of cellulose bio mass that makes it such a challenge to breakdown into simple sugars that can be converted to ethanol.

A current barrier to cellulose ethanol production is lower sugar yield. What is required is more effective pre treatment to solubilize hemi cellulose and cellulose which are locked into a rigid cell-wall structure by lignin. Use of harsh thermo-chemical pretreatments generate chemical by-products that inhibit enzyme hydrolysis and decrease the productivity of fermentative microbes. The crystalline structure of cellulose makes it more difficult for aqueous solutions of enzymes to convert cellulose to glucose.

SMC circumvents this barrier to higher sugar yield with high speed water jets resulting from ultrasonic cavitation bubble collapse which break open and pulverize the lignin-cellulose crystalline casing thereby exposing the cellulose and hemi cellulose molecules. The associated temperature of 5,000° K. and pressure of 500 atmospheres initiates flameless combustion of these cellulose molecule atomic structures which by dissociation converts cellulose to glucose.

In the earlier referenced experiments, with the onset of SMC fish food mineralization (dissociation), the presence of lignin became apparent when the transparent aqueous medium was progressively dyed dark brown. However, by the end of SMC mineralization and commencement of nitrification the aqueous medium had returned to its original transparent state. This confirmed that SMC dissociation had eliminated the lignin dye residue.

Environmental Impact:

Sono-Molecular-Conversion of orthophosphoric acid (H₃PO₄) reduces it to the phosphate anion (PO₄) effluent discharge into streams, rivers, lakes and estuaries to natural occurring levels and well below regulatory standards.

In the year 2005, U.S. Steel's ammonia discharge rate into Lake Michigan was 19 lbs/day, British Petroleum's 2007 Permit allows 1582 lbs/day, and unregulated paper makers discharge approximately 61,000 lbs/day.

In a sono-molecular conversion system, aqueous entrained gases such as nitrogen (N₂) and ammonia (NH₃, if present) are rapidly released to atmosphere with a jet pump venturi faucet which prevents these entrained gases from being discharged into public waterways or large lakes. The jet pump venturi faucet device features a high vacuum (⅓ atmosphere) rather than the design-limited low vacuum ( 1/100 atmosphere) illustrated and claimed in U.S. Pat. No. 5,665,141.

The sono-molecular conversion ultrasonically pulverizes low-level concentration (ppm) suspended organic solids into micron size inorganic particles, thereby posing no sludge-forming organic solids ecosystem threat to public waterways or large lakes.

Sono-molecular conversion, due to the extreme pressures and temperatures involved in ultrasonic transient cavitations, concurrently destroys bacteria, viruses, algae, parasites, and converts PCB and DDT into harmless short term acids. It has also been shown to effect cold evaporation of methyl mercury for filter collection before detoxified effluent is returned into the cleaning tanks.

A battery of bio-film SBRs' removing 74,920 lb of ammonia would emit 138 tons of CO₂ into the stratosphere. By contrast; one sono-molecular conversion system removing 74,920 lb of ammonia emits no green house gases.

Sono-molecular conversion reduces PCB and DDT into harmless short-term acids and has the potential to effect cold evaporation of methyl mercury for collection. An SBR bio-film has no impact on these industrial pollutants of the Great Lakes eco system.

Sono-molecular conversion converts organic waste to inorganic and destroys algae and parasites that pollute the Great Lakes eco system. SBR bio-film has no impact on these pollutants.

Carbon Dioxide:

The same structure disclosed herein used for treating ammonia, nitrites, and nitrates, can also be used to reduce CO₂ content in waste water. CO₂ in passing through sono-molecular-conversion at 5000° K. and 500 atmospheres undergoes thermal/pressure decomposition and subsequent dissociation to CO₂, CO+O₂. After dissociation, 222.3 kg of CO₂ yields 72.69 kg CO₂+95.16 kg CO+54.48 kg O₂. Since CO₂ and CO gases are continuously discharged to atmosphere there will be no build-up.

Although the invention has been described in terms of particular embodiments and applications, one of ordinary skill in the art, in the light of this teaching, can generate additional embodiments and modifications without departing from the spirit of or exceeding the scope of the claimed invention. Accordingly, it is to be understood that the drawings and the descriptions herein proffered by way of example to facilitate comprehension of the invention and should not be construed to limit the scope thereof. 

1. A sono-molecular-conversion method for treating waste water, the method comprising: (a) feeding the waste water containing organic matter through a first sono-molecular conversion device including a plurality of ultrasound transducers; (b) applying ultrasonic energy to the waste water containing the organic matter by the sono-molecular conversion device to ultrasonically collapse microsized bubbles with transient cavitation in said waste water containing organic matter to effect mineralization of the organic matter into ammonia therein by sono-molecular-conversion; (c) feeding the waste water containing the ammonia through a second sono-molecular conversion device including a plurality of ultrasound transducers; and (d) applying ultrasonic energy to the waste water containing the ammonia by the sono-molecular conversion device to ultrasonically collapse microsized bubbles with transient cavitation in said waste water containing the ammonia to effect nitrification of the ammonia into nitrates and nitrites therein by sono-molecular-conversion.
 2. The sono-molecular-conversion method according to claim 1, further comprising: feeding the waste water containing organic matter through a settling tank prior to passing the waste water containing organic matter to the first sono-molecular conversion device.
 3. The sono-molecular-conversion method according to claim 2, further comprising: feeding the waste water containing organic matter through a degritter prior to passing the waste water containing organic matter to the first sono-molecular conversion device.
 4. The sono-molecular-conversion method according to claim 2, further comprising: feeding some of the waste water from the settling tank into the second sono-molecular conversion device without having it pass through the first sono-molecular conversion device.
 5. The sono-molecular-conversion method according to claim 1, further comprising: feeding the waste water containing organic matter through a degritter prior to passing the waste water containing organic matter to the first sono-molecular conversion device.
 6. The method according to claim 1, wherein the method further includes continually or periodically monitoring the ammonia levels and automatically adjusting the intensity of the ultrasonic energy in response to changes in the ammonia levels.
 7. The method according to claim 1, wherein the method further includes continually or periodically monitoring the nitrites and nitrates levels and automatically adjusting the intensity of the ultrasonic energy in response to changes in the nitrites and nitrates levels.
 8. The method according to claim 1, wherein the sono-molecular conversion device comprises: a primary chamber having a first maximum diameter; a first conduit leading into a first end of the primary chamber; a second conduit leading into a second end of the primary chamber, wherein the first end is at an opposite side of the primary chamber as the second end; and a plurality of ultrasound transducers arranged at the second end of the primary chamber so as to emit ultrasonic energy into the primary chamber.
 9. The method according to claim 8, wherein the plurality of ultrasound transducers are focused at the first end of the chamber.
 10. The method according to claim 9, wherein a diameter of each of the first and second conduits is smaller than the first maximum diameter of the primary chamber.
 11. The method according to claim 9, wherein a velocity of the water is highest in the first and second conduits than in the primary chamber.
 12. The method according to claim 11, wherein a pressure of the water is lowest in the first and second conduits than in the primary chamber. 